Ibuprofen: Clinical Pharmacology, Medical Uses and Adverse by Wilton C. Carter, Brant R. Brown

By Wilton C. Carter, Brant R. Brown

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Table 3. S. S. S. Ref. 7 [165] [92] [46] [48] [47] [49] [156] [156] Values indicated alone are mean values (maximum values). LOQ: limit of quantification. LOD: limit of detection. : not detected. AC: activated carbon GAC: granular activated carbon. *(mg day -11000 inh-1). **(g d-11000 inh-1). A preliminary analysis of ibuprofen removal efficiencies achieved by different water treatments can be obtained from the data gathered in Table 3. Around 60 % of STPs and WWTPs use primary treatment followed by secondary biologic treatment with activated sludge, and the removal efficiencies range from values as low as 20 % [86, 93] to the complete removal [73, 110, 123].

In spite of the sizeable amounts of human drugs released to the environment (see Tables 2, 3 and 4), concise regulations for ecological risk assessment are largely missing. Only in the last few years, regulatory agencies have issued detailed guidelines on how pharmaceuticals should be assessed for possible unwanted effects on the environment. The first requirement for ecotoxicity testing, as a prerequisite for registration of pharmaceuticals, was established in 1995, according to the European Union (EU) Directive 92/18 EEC and the corresponding “Note for Guidance” [162] for veterinary pharmaceuticals.

Changes in seasonal temperature patterns are also a critical factor in constructed wetlands efficacy [199, 220, 232]. In fact, temperature appears to be one of the most determinant parameters in PPCPs biodegradation, as nitrifying and proteolitic bacteria living in constructed wetlands, usually reach their optimal activity at 15 – 25 °C [238]. Once ibuprofen removal in wetland follows mostly a biodegradation pathway, higher removals are observed at summer conditions (see Table 7). The work published by Hijosa-Valsero et al.

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